Removal of radioactive materials and heavy metals from water using magnetic resin

ABSTRACT

Magnetic polymer resins capable of efficient removal of actinides and heavy metals from contaminated water are disclosed together with methods for making, using, and regenerating them. The resins comprise polyamine-epichlorohydrin resin beads with ferrites attached to the surfaces of the beads. Markedly improved water decontamination is demonstrated using these magnetic polymer resins of the invention in the presence of a magnetic field, as compared with water decontamination methods employing ordinary ion exchange resins or ferrites taken separately.

The United States Government has rights in this invention pursuant toContract No. DE-AC04-76DP03533 between the United States Department ofEnergy and Rockwell International Corporation.

BACKGROUND OF THE INVENTION

This invention relates generally to decontamination of water, and moreparticularly, to a method for removing heavy metals and actinides fromcontaminated water using a magnetic polymer resin, a method forpreparation of the resin, the resin itself, and a method forregenerating and reusing the magnetic polymer resin.

Wastes generated by government and industry as a result of the nuclearfuel cycle, nuclear weapons development and production and otherindustrial processes commonly include water contaminated with variousheavy metals and radioactive materials including measurable amounts ofactinides. Water decontamination methods available presently fall intotwo basic types: 1) maximum dilution, and 2) maximum concentration andsubsequent removal of the contaminant. Maximum dilution achievesdecontamination by dramatically increasing the amount of otherwise inertmaterials in a contaminated water sample and effectively decreasingcontaminant concentration prior to either storage or disposal by releaseinto the environment. Maximum concentration and removal, on the otherhand, typically involves water purification methods includingadsorption, ion exchange, chemical precipitation, flocculation,filtration and biological retention. Such purification methods allow forthe concentration and removal of contaminants in order that thecontaminants may be stored or disposed of in isolated hazardous wasterepositories. Varieties of these methods have been used in managingradioactive wastes, nonradioactive wastes and mixed wastes. The presentinvention involves concentration and removal of contaminants.

It has been demonstrated that mixed valence iron oxide compounds, orferrites, are effective in removing heavy metals and suspended solidsfrom aqueous media. Due to their unique chemical structure, ferrites maycontain one or more iron atoms capable of being replaced by other metalions. This characteristic, together with ferrites' strongly magneticcharacter, make them particularly suited to applications associated withwaste water decontamination. Toshio Takada, "Removal of Heavy Metal Ionsfrom Waste Water by Ferritization," Koga to Taisaku 13, 37 (1977);Toshiyuki Iguchi, Toyokazu Kamura, and Masahiro Inoue, "Ferrite Processfor Treatment of Waste Water Containing Heavy Metals," Poll. Prev. andDev. Tech. 10, 49 (1979); Tomio Nagashima, "Removal of Hazardous Metalsfrom Waste Water," Japan, Kokai 77 77,465 (1977); Masakatu Sano,"Removal of Hazardous Metals from Waste Water," Japan, Kokai 77 67,156(1977); Izuru Sugano, "Removal of Hazardous Metals from Waste Water,"Japan, Kokai 77 67,154 (1977); Christopher de Latour and Henry Kolm,"Magnetic Separation in Waste Water Pollution Control," IEEE Trans. onMagnetics 11, 1570 (1975). Magnetite, a common ferrite, is a strongadsorbent which has been used successfully for removing organicmaterials and biological matter such as algae, bacteria, viruses, andseeds from water. Thomas E. Boyd, M. J. Cusick, and James D. Navratil,"Ferrite Separation Science and Technology," Recent Developments inSeparation Science, 8, pp. 207-232, N. N. Li and J. D. Navratil, Eds.,CRC Press, 1986.

Ferrites have also been demonstrated to be effective in removal ofactinides (thorium, uranium, plutonium and americium) from waste watergenerated at the nation's nuclear weapons production facilities. Ferriteremoval of actinides can be accomplished using several differenttechniques including mixing prepared ferrites with aqueous wastes andpreparing ferrites in situ in waste solutions. "Removal of RadioactiveMaterials from Waste Solutions Via Magnetic Ferrites," Thomas E. Boyd,Robert L. Kochen, and Marlene Y. Price, ANS Topical Meeting on Treatmentand Handling of Radioactive Wastes, Richland, Wash. (1982); Robert. L.Kochen, "Actinide Removal From Aqueous Solution with ActivatedMagnetite," RFP-4100, Rockwell International, Rocky Flats Plant, Golden,Colo. (1987); Thomas E. Boyd, Robert L. Kochen, "Ferrite Treatment ofActinide Waste Solutions: Continuous Processing of Rocky Flats ProcessWaste," RFP-3476, Rockwell International, Rocky Flats Plant, Golden,Colo. (1983), Thomas E. Boyd, Robert L. Kochen, James D. Navratil andMarlene Y. Price, "Actinide Aqueous Waste Treatment Studies UsingFerrites," Radioactive Waste Management and the Nuclear Fuel Cycle,4(2), 1983.

A different approach to waste water decontamination involves the use ofanion exchange resins for the removal of various contaminants fromaqueous media. Polyamine-epichlorohydrin-type resins were firstdemonstrated to be effective weakly basic anion exchange resinsapproximately thirty years ago. C. A. Feldt and G. T. Kekish, "WeaklyBasic Anion Exchange Resins," U.S. Pat. No. 3,092,617 (1963). Organicion exchange resins are commonly used in chemical treatment ofcontaminated water in both industrial waste water treatment and generalwater resources engineering. Extensive research efforts have been madeto develop organic ion exchange resins that are suited to adsorbingparticular organic and inorganic contaminants. Alone, however, organicion exchange resins are not especially effective for purposes ofremoving actinides from water, especially since noncharged polymericspecies can be present in the water.

Due to the fact that large amounts of waste water containing heavymetals, or actinides, or both, are being generated, stored and disposedof in the United States and elsewhere, improved methods for handling anddecontaminating such waste water are needed. The present invention helpsto serve this need by providing a highly effective means for removingheavy metals and actinides from water.

SUMMARY OF THE INVENTION

The described invention greatly enhances removal of actinide and heavymetal contaminants from water as compared with existing waterdecontamination processes. By joining magnetic ferrites with polymerresins to produce magnetic ion exchange resins, and by utilizing theresins in the presence of a magnetic field, the invention yieldsmarkedly improved decontamination results due to an apparent andunexpected synergism between the individual mechanisms associated withferrite decontamination systems, ion exchange resins and an externalmagnetic field.

Accordingly, it is an object of the present invention to provide amethod for decontamination of wastes containing water and heavy metals(including, but not limited to cobalt, copper, arsenic, chromium,silver, lead, mercury, and cadmium, and combinations of those metals),beryllium, or actinides, or a combination of them which utilizesmagnetic ferrites, anion exchange resins, and a magnetic field incombination.

It is another object of the invention to provide a method which exploitsthe apparent synergism between magnetic ferrites, anion exchange resins,and a magnetic field for purposes of contaminant removal from water.

It is yet another object of the invention to provide a method forpreparation of magnetic ion exchange resins.

It is yet another object of the invention to enhance of thedecontamination effect by carrying out the method in the presence of amagnetic field.

It is yet another object of the invention to provide magnetic ionexchange resin polymers, themselves.

It is yet another object of the invention to provide a method forregeneration and reuse of spent magnetic polymers.

It is yet another object of the invention to enhance the regeneration ofspent magnetic polymers by carrying out the regeneration step outside ofthe presence of the magnetic field.

Additional objects, advantages and novel features of the invention willbecome apparent to those skilled in the art upon examination of thefollowing description or may be learned by practice of the invention.The objects and advantages of the invention may be realized and attainedby means of the methods, instrumentalities and combinations particularlydescribed in the appended claims.

The foregoing objects and others are accomplished in accordance with thepresent invention by providing a weak-basepolyamine-epichlorohydrin-type anion exchange resin beads with ferriteparticles such as magnetite attached to outer bead surfaces. This resinis synthesized by crosslinking polyethyleneimine withammonia-epichlorohydrin polymer under suspension conditions with asurfactant and an activated magnetite. The result is a magneticpolyamine-epichlorohydrin resin that exhibits good flow-throughproperties when used in a column mode in the presence of a magneticfield and provides an effective means for removing both heavy metalcontaminants and actinides from water. The objects are also accomplishedby providing methods for preparation, use, regeneration and reuse ofsuch a resin as set forth in detail throughout the remainder of thisdisclosure.

BRIEF DESCRIPTION OF THE DRAWINGS

FIG. 1(a) is a photomicrograph of magnetic polyamine-epichlorohydrinresin beads ranging in size from <0.125 to 0.063 mm taken at 50×magnification.

FIG. 1(b) is a photomicrograph of magnetic polyamine-epichlorohydrinresin beads ranging in size from <0.125 to 0.063 mm taken at 500×magnification.

FIG. 1(c) is a photomicrograph of magnetic polyamine-epichlorohydrinresin beads ranging in size from <0.125 to 0.063 mm taken at 200×magnification.

FIG. 1(d) is an iron print of magnetic polyamine-epichlorohydrin resinbeads ranging in size from <0.125 to 0.063 mm taken at 200×magnification.

FIG. 2 shows a schematic drawing of an apparatus preferred for thedecontamination method of the invention.

FIG. 3 is a graphic representation of results obtained for plutoniumremoval using the invention.

FIG. 4 is a graphic representation of results obtained for americiumremoval using the invention.

FIG. 5 is a graphic representation comparing results obtained forplutonium removal using magnetic polyamine-epichlorohydrin resin in thepresence of a magnetic field versus plutonium removal using the resin inthe absence of a magnetic field.

FIG. 6 is a graphic representation comparing results obtained forplutonium removal using magnetic polyamine-epichlorohydrin resin in thepresence of a magnetic field versus using non-magnetic polyamineepichlorohydrin resin.

DETAILED DISCUSSION

Significantly enhanced decontamination of water is achieved where ionexchange materials or sorbents are improved by attaching magneticferrites to the surfaces of the ion exchangers. A wide variety ofmagnetic ferrites having the formula MO.M₂ O₃ may be used. In this case,one M is iron and the other M may be iron, barium, magnesium, calcium orother similar elements. The ion exchangers to which the magneticferrites are attached, may include anion or cation exchange polymers,inorganic ion exchangers, sorbents or other materials, such as glasswool, sea sand and the like, which are capable of adsorbing watercontaminants and supporting the ferrites. In the preferred embodiment,polyamine-epichlorohydrin resin beads are synthesized with magnetiteparticles attached to the outer surfaces of the beads.

FIGS. 1(a) through 1(d) illustrate the size and shape of magneticpolyamine-epichlorohydrin (MPE) beads synthesized using the process ofthis invention. Also shown are iron prints taken of MPE beads depictingthe distribution of ferrite particles over the surfaces of the beads.The beads depicted in FIGS. 1(a) through 1(d) range in size from 0.063mm to just less than 0.125 mm in diameter, however, larger and smallerbeads can also be synthesized. A significant advantage associated withthese ferrite-coated beads lies in their large surface areas whichpermits efficient contact between magnetite-embedded resin andcontaminated water as it is pumped through the column. The size of beadsselected for a particular application depends on desired surface areaand flow-through characteristics.

The polyamine-epichlorohydrin resin beads with attached ferriteparticles are synthesized using a two-step process. First,epichlorohydrin is slowly added to a stirred aqueous ammonia solutionthus promoting an exothermic reaction which yields a clear, transparentammonia-epichlorohydrin polymer. Following the reaction, this polymer isallowed to cool to ambient temperature.

In the second step, the ammonia-epichlorohydrin polymer is combined withpolyethyleneimine (10% aqueous solution) and activated ferrite in aflask containing toluene and a surfactant. This mixture is then stirredat elevated temperature while the azeotropic mixture of water andtoluene are refluxed for a period of several hours until magneticpolyamine epichlorohydrin (MPE) resin is produced. The resulting beadsmay be filtered out of the liquid medium, and then dried and sortedaccording to size.

Non-magnetic polyamine-epichlorohydrin (PE) resin can also besynthesized using the same procedure, except that no ferrites are addedin the second step. PE resin was synthesized in connection with theexperiments described below for the purpose of demonstrating theapparent synergism between ferrites in a magnetic field andpolyamine-epichlorohydrin resin for purposes of water decontamination.

FIG. 2 illustrates the preferred apparatus for practicing the invention.This experimental set-up was used in the examples that follow. Accordingto the preferred embodiment, a vertical glass column (1) is placedbetween the pole faces (2a) and (2b) of an electromagnet. A piece ofstainless steel wool (3) is positioned inside the column, approximatelyequidistant from both ends, to provide a barrier which is penetrable byliquid, but which is substantially impenetrable to solid beads. At thebottom of the column is positioned a stopcock (4) to which is attachedone end of a piece of inlet tubing (5). The opposite end of the inlettubing is placed in operative association with a pump means (6) which,in turn, is inoperative association with a feeder tube (7) leading toand terminating in a source container (8) bearing contaminated solution.The arrangement of the feeder tube, pump means, and inlet tube isvariable according to the type of pump means used. It is necessary onlyto be able to pump solution from a source container into and through theglass column.

Another section of tubing, an effluent tube (11), is adjoined to the topof the glass column and terminates in an effluent container (9) intowhich decontaminated solution is permitted to flow. Finally, magneticpolyamine-epichlorohydrin (MPE) resin beads (10) are emplaced in thecolumn above the stopcock and below the stainless steel wool.

According to the preferred method of the invention, MPE resin beads areactivated with barium hydroxide and slurried with NaOH solution so as toachieve pH of 12.0. Pretreatment (or activation) of the magnetitesurface with hydroxyl ions greatly influences the extent to which themagnetite acts as an actinide adsorbent. Magnetite activated with bariumhydroxide is effective over a pH range of 11.0 through 13.5 and lowersplutonium concentrations from 10⁻⁴ to 10⁻⁸ grams per liter. Similarly,sodium hydroxide-activated magnetite lowers plutonium concentrations inwater from 10⁻⁴ to 10⁻⁸ grams per liter at pH 12 to 13.

The resin bead slurry is then pumped upward into the column while amagnetic field is applied with the electromagnet. When waste solution isnot being actively decontaminated and the pump is turned off, thestopcock may be closed to prevent MPE beads from passing out of thebottom of the column.

With the column thus prepared, the stopcock is opened and aqueoussolution contaminated with actinides, heavy metals, or both, is pumpedinto the bottom of the column, and through the slurry of MPE beads. Amagnetic field is constantly applied using the electromagnet. As thesolution is pumped through the resin bead slurry in the presence of themagnetic field, heavy metal and actinide contaminants adsorb onto thebeads. Liquid thus decontaminated then passes upward out of the column,through the effluent tube and into the effluent container.

The mechanism of the adsorption process is complex. Fundamentally,however, the adsorption of cations increases with pH, as the negativecharge on the magnetite increases above the isoelectric point of 6.9. D.R. Dixon, Interaction of Alkaline-Earth-Metal Ions With Magnetite,Colloids and Surfaces, 13, pp 273-286, 1985. The isoelectric point isthe pH at which the positive and negative charges on the molecule arebalanced, and the molecule does not move in either direction when placedin an electric field. When pH is lowered below the isoelectric point,the surface charge on the magnetite becomes positive and the cations arereleased.

After the MPE beads adsorb the contaminants, they can be cleaned andreused. In regeneration, the surface charge on the magnetite can be madepositive (for cation release) by treating with mineral acid. Both nitricacid (0.1M and 3.0M) and hydrochloric acid (0.1M and 3.0M) wereevaluated for removing actinide activity from MPE resin. The 3.0M HClwas the more effective solution for removing the actinide activity.Removal of the actinides in this fashion from the MPE resin requiresthat the magnetite be completely dissolved from the resin matrix.

In the preferred embodiment, cleaning of the beads is effected bywashing heavy metal and actinide contaminants off of them using eitherKOH or NaOH at a pH greater than 12.5. MPE beads reactivated in thismanner can be reslurried and used again in the same fashion that theywere used originally. Besides KOH and NaOH, aqueous solutions ofcomplexing agents, such as EDTA, citrate, and the like, may also be usedfor elution of the beads.

The decontamination process of the invention may be used to removeberyllium and a wide variety of heavy metals (including cobalt, copper,arsenic, cadmium, silver lead, mercury and cadmium) from aqueous waste.Likewise, actinides such as thorium, uranium, plutonium, americium andothers can be effectively removed from aqueous solutions according tothis invention. Combinations of these elements can likewise be removed.

Actinide decontamination results are depicted in FIGS. 3, 4, 5 and 6.FIG. 3 shows the results of an experiment in which approximately 350liters of plutonium-contaminated water were passed through a column suchas is described above. The initial plutonium concentration in thecontaminated water prior to treatment was 1.28×10⁻⁴ grams Pu-239 perliter and the MPE resin bead size ranged from less than 0.125 mm indiameter to 0.063 mm in diameter. The flow rate upward through thecolumn was 3.5 ml/min./cm² (0.87 GPM/Ft²) with 0.3 Tesla applied to theelectromagnet. (It is noted here that varying degrees of decontaminationcan be accomplished using any field strength within the range of 0.2 to1.0 Tesla.) The technique by which the MPE resin beads were synthesizedis described below in Example 1. For purposes of collecting these data,column effluent was collected in 250 ml aliquots and analyzed foractinide concentration at one-liter intervals. After 270 liters ofsolution were processed, the effluent was collected in one-literaliquots and analyzed for actinide concentration at five-literintervals.

The graph in FIG. 3 shows that the amount of plutonium in the effluentwater decreased dramatically at the outset as contaminated water passedthrough the matrix of MPE resin beads. This indicates that most of theplutonium present in the contaminated water had been trapped by the MPEbeads. Only after the beads started to become saturated did theconcentration of plutonium in the effluent start to rise. Using theinvention, plutonium concentrations in 325 liters of water were loweredfrom 1.28×10⁴ - g/l to 2.77×10⁻⁸ g/l with 20 grams of MPE resin.

FIG. 4 shows results similar to those depicted in FIG. 3, except thatthey pertain to the rate of americium removal by MPE resin beads wherethe initial americium concentration in the water prior to treatment was3.57×10⁻⁷ grams Am-241 per liter. The remainder of the parameters andthe sampling regimen were the same as those stated above for FIG. 3.Again, very low effluent concentrations of americium were detected untilthe MPE beads started to become saturated. Using the invention,americium concentrations in 325 liters of water were lowered from3.57×10⁻⁷ g/l to 7.17×10⁻¹⁰ g/l with 20 grams of MPE resin.

FIG. 5 shows the results of a run wherein MPE resin beads ranging indiameter from less than 0.125 mm to 0.063 mm reduced plutoniumconcentration in water steadily from approximately 10⁻⁴ g/l to nearly10⁻⁸ g/l in the presence of a magnetic field with a field strength ofabout 0.3 Tesla. However, when the magnetic field was removed, theefficacy of the plutonium removal by the MPE beads declineddramatically.

Similarly, FIG. 6 shows the enhanced plutonium removal capability of MPEin comparison with non-magnetic polyamine-epichlorohydrin resin (PE) inthe presence of a magnetic field. In this run, both types of resin weretested for their capability of removing plutonium from contaminatedwater in the presence of a magnetic field with a field strength of about0.3 Tesla. Although there was an initial decrease in plutoniumconcentration with both types of resin, the capability of PE to removeplutonium diminished quickly. The MPE, on the other hand, reducedplutonium contamination to lower concentrations than did the PE, and theMPE remained effective for treating a significantly larger volume ofplutonium contaminated water.

Ferrites alone can also be used to remove actinides from water, althoughthey are less effective than MPE in the presence of a magnetic field.Using the invention, 8,600 liters of actinide-contaminated water can besuccessfully treated with one liter of MPE resin. (The density of wetMPE resin is 0.53 g/cm³.) Two grams of magnetite are required to treatone liter of waste water by lowering plutonium concentration from 10⁻⁴g/l to 10⁻⁸ g/l. Thomas E. Boyd and Robert L. Kochen, "Ferrite treatmentof Actinide Waste Solutions: Continuous processing of Rocky FlatsProcess Waste," RFP-3476, Rockwell International, Rocky Flats Plant,Golden Colo., Mar. 18, 1983. Typically, therefore, 650 grams ofactivated magnetite would be required to lower plutonium concentrationin 325 liters of water from 10⁻⁴ g/l to 10⁻⁸ g/l. Similar results havebeen demonstrated with only 20 grams of MPE resin.

The present invention's capability of highly effective removal ofactinides depends on an apparent synergistic effect involving thecombination of both polyamine-epichlorohydrin resin and ferrites in thepresence of a magnetic field. Neither PE resin alone nor ferrites alonecan achieve comparable results given similar conditions.

Without further elaboration, it is believed that one skilled in the artcan, using the preceding description, utilize the present invention toits fullest extent. The following examples are to be construed as merelyillustrative and not limitative of the remainder of the disclosure inany way whatsoever.

EXAMPLE 1

Resin Preparation: Polyamine-epichlorohydrin resin beads are synthesizedwith ferrite particles attached to the outer bead surfaces. First, 1.7moles (103 g) of aqueous ammonia solution (28% ) are placed into aone-liter three-necked flask. The flask is equipped with a mechanicalstirrer, a thermometer, and a 125-ml dropping funnel. One mole (92.5 g)of epichlorohydrin is added by drops through the dropping funnel to theaqueous ammonia solution being stirred at 500 rpm. The epichlorohydrinis added over a one-hour period with the rate of addition sufficient tomaintain an exothermic reaction temperature of 90°±2° C. At the end ofthe one-hour period, a clear, transparent polymer(ammonia-epichlorohydrin) is removed and cooled to ambient temperature(23°±2° C).

Next, 95.0 g of previously prepared ammonium-epichlorohydrin polymer,58.0 g polyethyleneimine (10% aqueous solution), and 9.0 g of wet,activated ferrite (in this case, magnetite) are added to a one-literthree-necked flask that contains 150 ml of toluene and 4.5 g Aerosol™GPG surfactant. The flask is equipped with a heating mantel, athermometer, a mechanical stirrer, a Friedrichs™ condenser (350-mm), anda Barrett™ water trap (20-ml).

Then, the mixture is stirred for five minutes at 1700 rpm and anadditional 5 g of epichlorohydrin is added to the flask. The temperatureis raised to 85°±2° C. and the mixture is then allowed to stir at 1000rpm while an azeotropic mixture of water and toluene are refluxed.Additional toluene (about 350 ml) is added as needed to allow therefluxing to continue. The refluxing is sustained for 4.5 hours and thewater is removed as necessary from the Barrett™ trap. At the end of theheating period, the product, a magnetic polyamine-epichlorohydrin resin,is cooled, filtered through Whatman™ No. 41 (20-25 micron) filter paper,air dried and sieved.

EXAMPLE 2

Column preparation: The upper portion of a glass chromatographic column(19 mm i.d×25 cm) is packed with a 10 cm plug of fine, No. 431 stainlesssteel wool. The column is then placed between the poles of anelectromagnet such that the bottom portion of the steel wool plug ispositioned amid the two poles. (Glass wool can be used in place of thestainless steel wool.) The bottom of the column is fitted with astopcock and the top of the column is fitted with a rubber stopper andexit tube. Tygon™ tubing is attached to both ends of the column.

Next, the magnetic polyamine-epichlorohydrin (MPE) resin is activated bystirring it with a solution of barium hydroxide (2.6 mmol per gram ofmagnetite) for 10 minutes at ambient temperature. The excess bariumhydroxide solution is then decanted and sodium hydroxide solution (pH12.0) is added to the wet MPE resin. This MPE slurry is then pumped(up-flow at 10 ml per minute via a peristaltic pump) into the glasscolumn while a field strength of 0.3 Tesla (3,000 Gauss) is applied bythe electromagnet. This results in a high-gradient magnetic effect thatis responsible for the high efficiency removal of heavy metal andactinide ions from the water. The magnetic field also helps to ensurethat the magnetic resin remains in the column while fluid is allowed toflow through.

We claim:
 1. An adsorptive process for removing contaminants from watercomprising the steps of:placing water contaminated with cationic speciesincluding actinides in contact with a magnetic polymer composition inthe presence of an external magnetic field, said magnetic polymercomposition comprising an anion exchange resin combined with magneticparticles, and permitting said cationic species to adsorb to saidmagnetic polymer composition.
 2. The method of claim 1 wherein saidcontaminants further include heavy metals.
 3. The method of claim 2wherein said heavy metals are selected from the group consisting of,cobalt, copper, arsenic, chromium, silver, lead, mercury, cadmium andany combinations of those elements.
 4. The method of claim 1 whereinsaid anion exchange resin comprises polyamine epichlorohydrin.
 5. Themethod of claim 1 wherein said magnetic particles comprise ferrite. 6.The method of claim 5 wherein said ferrite is magnetite.
 7. The methodof claim 1 wherein said magnetic polymer substance comprises weak-basepolyamine epichlorohydrin anion exchange resin beads with ferriteparticles attached to the outer surfaces of said beads.
 8. The method ofclaim 1 wherein said magnetic polymer substance comprises weak-basepolyamine epichlorohydrin anion exchange resin beads with ferriteparticles attached to the outer surfaces of said beads and wherein saidbeads are synthesized by crosslinking polyethyleneimine with ammoniaepichlorohydrin polymer under suspension conditions in the presence of asurfactant and an activated magnetite.
 9. The method of claim 1 furthercomprising the steps of:placing said magnetic polymer substance inside avertical column; placing said vertical column between the poles of amagnet; and pumping said contaminated water upward through said columnwhereby said contaminated water experiences contact with said magneticpolymer substance in the presence of a magnetic field.
 10. The method ofclaim 9 wherein said magnetic polymer substance is a magnetic polyamineepichlorohydrin resin.
 11. The method of claim 10 wherein said magnet isan electromagnet which exerts a magnetic field with a strength withinthe range of about 0.2 to 1.0 Tesla.
 12. The method of claim 10 whereinsaid magnet is an electromagnet which exerts a magnetic field with astrength of about 0.3 Tesla.
 13. The method of claim 1 wherein saidcontaminants include beryllium and heavy metals.
 14. The method of claim13 wherein said heavy metals are selected from the group consisting ofcobalt, copper, arsenic, chromium, silver, lead, mercury, cadmium andany combinations of those elements.
 15. The method of claim 1 whereinsaid contaminants further include beryllium.
 16. A method fordecontaminating water containing actinides comprising the stepsof:combining magnetic polyamine-epichlorohydrin resin with bariumhydroxide to form activated magnetic polyamine-epichlorohydrin resin;decanting any excess barium hydroxide from said activated magneticpolyamine-epichlorohydrin resin; adding sufficient sodium hydroxide tosaid magnetic polyamine-epichlorohydrin resin to yield a magneticpolyamine-epichlorohydrin slurry having a pH of about 12.0; placing saidslurry into a vertical column bearing a liquid penetrable barrierlocated inside said column, approximately equidistant from both ends ofsaid column; placing said column between the poles of an electromagnetsuch that said slurry is located between said poles; applying to saidslurry an electromagnetic field with a field strength of about 0.3Tesla; and pumping contaminated water containing actinides upwardthrough said slurry within said column.